Porewater-Derived Blue Carbon Outwelling and Greenhouse Gas Emissions in a Subtropical Multi-Species Saltmarsh

1 Introduction

Vegetated saltmarshes are crucial coastal blue carbon ecosystems with high carbon stocks and sequestration (McLeod et al., 2011). Atmospheric CO₂ photosynthetically sequestered via saltmarsh vegetation can be stored in biomass and then buried in sediments (Duarte et al., 2005; Lo Iacono et al., 2008). Although saltmarshes and other coastal wetlands, such as mangroves and seagrasses, cover only 0.2% of the global ocean surface, 50% of the carbon burial in ocean sediments originates from these coastal wetlands (Duarte et al., 2013). While saltmarshes are considered an important carbon sink, sediment carbon would potentially release from soil (Herrmann et al., 2015; Najjar et al., 2018). Microorganisms can cause decomposition of some sediment carbon into greenhouse gases (e.g., CO₂ and CH₄) and organic/inorganic carbon matter (Tang et al., 2018; Chen et al., 2020b). Then, these decomposed carbon species can be partially released into the adjacent ocean through porewater exchange (Santos et al., 2019; Liu et al., 2021; Tamborski et al., 2021; Chen et al., 2022; He et al., 2022). Globally, considerable amounts of carbon were transported into coastal waters through mangrove groundwater flow, which accounts for 29–48% of global riverine export to the ocean (Chen et al., 2018). However, limited studies focus on porewater-derived carbon exports and greenhouse gas emissions in saltmarsh ecosystems.

The flow of water through continental and insular margins, from the seabed to the coastal ocean, was defined as submarine groundwater discharge (Taniguchi et al., 2019). In saltmarshes, submarine groundwater discharge mainly relates to processes with sub-meter length scale (i.e., tidal and wave pumping, shear flow, and ripple migration), which can be more specific to porewater exchange (Taniguchi et al., 2019; Garcia-Orellana et al., 2021). As the surface water-groundwater exchange in coastal wetlands is mainly seawater circulation rather than fresh groundwater discharge, to emphasize the seawater circulation process in the root zone of coastal wetlands, the surface water-groundwater exchange is usually expressed by porewater exchange (e.g., Tait et al., 2016; Santos et al., 2019; Chen et al., 2021b; Chen et al., 2022; Wang et al., 2022). The interaction between porewater/groundwater and surface water is significantly affected by bioturbations, such as crab burrows (Xin et al., 2009; Xiao et al., 2020; Santos et al., 2021b; Xin et al., 2022). Quantifying the porewater exchange rate is essential to determine the transportation of carbon species across the sediment-water interface. Radon (²²²Rn) is a useful natural radioisotope for quantifying carbon exports associated with porewater exchange by integrating ²²²Rn fluxes that occur within a broad area of influence (Correa et al., 2021). ²²²Rn has been employed to estimate porewater exchange rates and related carbon fluxes in mangroves (Chen et al., 2018; Taillardat et al., 2018; Chen et al., 2021a; Wu et al., 2021) and saltmarshes (Chen et al., 2021b; Correa et al., 2021; Liu et al., 2021).

Carbon burial rates in saltmarshes have been quantified 1–3 orders of magnitude higher than those in terrestrial forests (McLeod et al., 2011; Duarte et al., 2013). Saltmarshes provide habitats for a diversity of salt- and/or saturation-tolerant plant species with high productivity (Guimond and Tamborski, 2021). However, plant biomass varies with species; thus, succession and invasion of saltmarsh vegetation can directly affect carbon composition and content in sediments (Seyfferth et al., 2020). In 1979, Spartina alterniflora, originally North America, was introduced into China for sediment accumulation due to strong root systems (Gao et al., 2012) and then rapidly spread in the eastern Chinese coastal region (Gao et al., 2014). Previous studies have found that sediment carbon burial rates change with different vegetation cover, such as Scirpus mariqueter and Spartina alterniflora (Xia et al., 2019). However, the mechanism and extent of porewater-derived carbon outwelling and greenhouse gas emissions in multi-species saltmarshes remain unknown.

Here, we hypothesized that porewater exchange is the major driving force of carbon outwelling and greenhouse gas emissions in multi-species salt marshes. We investigated spatial ²²²Rn, carbon (dissolved inorganic carbon (DIC) and dissolved organic carbon (DOC)), and greenhouse gas (CO₂ and CH₄) distributions for both intertidal porewater and surface water in a subtropical multi-species saltmarsh (Andong Shoal, China). In addition, we analyzed the contents of organic carbon, nitrogen, and δ¹³C isotopes in different saltmarsh vegetation. The objectives of this study were to (1) trace the origin of organic carbon in saltmarsh sediments, surface water, and porewater using the δ¹³C carbon isotope signature; (2) quantify the porewater exchange rate using a ²²²Rn mass balance model; and (3) estimate the fluxes of porewater-derived carbon outwelling and greenhouse gas emissions.

2 Materials and Methods

2.1 Study Region

Field investigations were performed in a multi-species saltmarsh, Andong Shoal, located on the protruding section of the tidal shoal on the south bank of Hangzhou Bay, China (Figure 1). Andong Shoal is an alluvial coast and has a subtropical monsoon climate with a mean annual temperature of 17.1°C and mean annual rainfall of 1381 mm (Cao et al., 2020). It is formed by the accumulation of sediments from the Yangtze and Qiantang River (Wu et al., 2008). The intertidal zone of Andong Shoal is 7–8 km wide (Song et al., 2014), with a developed creek system due to macrotidal conditions (Li and Xie, 1993). An irregular semidiurnal tide exists in this region, with a mean tidal range of 5.5 m (Huang et al., 2020). The vegetation in the saltmarsh includes not only local species such as Scirpus mariqueter, Suaeda glauca, and Phragmites australis (C3 plant species), but also invasive species such as Spartina alterniflora (C4 plant species) (Wang et al., 2015).

Figure 1 (A) Location of the study area (Andong Shoal); (B) Sampling stations for creek surface water, sediments and vegetations.

2.2 Sampling and Analytical Methods

2.2.1 Surface Water and Porewater

Field work was performed in saltmarsh tidal creeks along the Andong Shoal (Figure 1) during the wet season (May 2021) due to its obvious porewater flow (Young et al., 2005; Chen et al., 2018). Surface water samples (n=36) were directly pumped into 2 L polyethylene bottles using the overflow method (Chen et al., 2018). Then, the sampling bottle was connected in a close air loop with a RAD-7 detector (Durridge) and a Picarro G4301 for measuring ²²²Rn and greenhouse gases (including CO₂ and CH₄), respectively (Santos et al., 2012). In addition, each water sample was filtered through 0.45-μm nylon filters into 60 mL polyethylene bottles without headspace, in triplicate for DIC/DOC, organic nitrogen, and stable carbon isotope (δ¹³C) measurements. These filtrates were preserved by a saturated HgCl₂ solution (Gatland et al., 2014; Santos et al., 2019), which can eliminate the influence on the amount of carbon species via the microorganism process. Surface water temperature, salinity, water depth, pH, and dissolved oxygen (DO) profiles were recorded using an EXO3 Multiparameter Sonde automated datalogger. Wind speed data was obtained from the China Meteorological Data Service Center (http://data.cma.cn/). To approach the ²²²Rn ingrowth from ²²⁶Ra, surface waters were slowly passed through MnO₂-impregnated acrylic fibers for ²²⁶Ra enrichment, and the fibers were then washed with Milli-Q water to remove slats and particles (Moore and Arnold, 1996). These ²²⁶Ra-enrichment fibers were sealed for three months and subsequently analyzed using a RAD-7 detector (Peterson et al., 2009).

Porewater bores (n=9) were installed along the saltmarsh creek to capture the spatial variability in the Andong Shole (Figure 1). Samples of porewater ²²²Rn, CO₂, and CH₄ were collected in 2-L polyethylene bottles and analyzed using the same methods as the surface water. The DIC/DOC, organic nitrogen, and δ¹³C samples were collected and treated as described earlier. In addition, the porewater temperature, salinity, pH, and DO were measured using a Multi 3430 WTW digital multi-parameter meter.

DIC and DOC samples of the surface water and porewater were analyzed using a TOC-L (Shimadzu, Japan) total organic carbon analyzer (Chen et al., 2018). DIC concentrations were directly measured by injecting water samples into the reactor with spiked hydrochloric acid. DOC concentrations were considered as the difference between the total dissolved carbon (TDC) and DIC. To determine the TDC concentrations, water samples were combusted in a 680°C tube with a catalyst. The measurement errors were ±4% for DIC and ±5% for TDC, with a precision of < ± 1%. Organic nitrogen represents the difference between total nitrogen and dissolved inorganic nitrogen (including NO₃-N, NO₂-N, NH₄-N). The concentrations of total nitrogen and dissolved inorganic nitrogen were measured using a San⁺⁺ continuous flow analyzer by adapting spectrophotometric method (Kroon, 1993; Liu et al., 2009). Organic ¹³C isotope samples were analyzed using an ISOPRIME100 (Elementar, Germany) stable isotope mass ratio spectrometer and calculated as δ¹³C values referring to the international standard Vienna Pee Dee Belemnite (VPDB) (Degens, 1969). Replicate analysis of the laboratory standard samples indicated a precision of ±0.16%.

2.2.2 Sediments and Saltmarsh Plants

Saltmarsh sediment samples were collected to estimate ²²²Rn diffusive flux using a sediment equilibration experiment (Corbett et al., 1998). One liter or 1.5 kg of sediment was incubated with 5 L of radium-free water in a sealed flask for three months. Once the dissolved ²²²Rn had equilibrated between water and sediment, 2 L of water was pumped into a polyethylene bottle, and the ²²²Rn concentration was analyzed using a RAD-7 detector. Sediment cores and saltmarsh plant samples, such as Scirpus mariqueter, Spartina alterniflora, Suaeda glauca, and Phragmites australis, were collected (Figure 1). The sediment samples were sealed in aluminum foil bags and stored at -40°C. For saltmarsh plants, each species was cleaned, separated into leaves, stems, and roots, and then stored using the same method as the sediment samples. Sediment and plant samples were analyzed for organic carbon, organic nitrogen, and δ¹³C values using a 253plus (Thermo Scientific, US) isotope ratio mass spectrometer (Pérez et al., 2020). The δ¹³C values were calculated by referring to the VPDB. The precisions were ±0.5% for organic carbon, ± 1% for organic nitrogen and ±0.05% for δ¹³C.

2.3 ²²²Rn Mass Balance Model, Carbon Outwelling and Greenhouse Gas Emissions

The ²²²Rn mass balance model (Burnett and Dulaiova, 2003) has been widely used to quantify advective porewater flux in saltmarshes and mangroves (e.g., Santos et al., 2019; Correa et al., 2021; Chen et al., 2022). The model integrates all ²²²Rn sources (e.g., imports from bay water during the flood tide, diffusion from sediments, and ingrowth from dissolved ²²⁶Ra) and sinks (exports during the ebb tide, atmospheric evasion, and radioactive decay). Surface water samples were collected during the highest tide level, because the sampling boat can reach the upstream sites at this time. Assuming all the creek water is discharged during ebb tide, the missing ²²²Rn represents porewater exchange in each tidal cycle. At steady state, integrating all of fluxes over a complete day, the porewater exchange flux (F_pw, Bq m^-2 d^-1) can be estimated as follows:

where ²²²Rn_sw is the average ²²²Rn activity (Bq m^-3) in surface water during the flood tide, Δv is the difference of water volume in creeks between high tide level and low tide level (m³ d^-1), F_atm is the ²²²Rn flux to the atmosphere (Bq m^-2 d^-1), which can be calculated by concentration gradients, wind speed and current (Chen et al., 2020a), λ is the ²²²Rn decay constant (0.182 d^-1), ²²²Rn_sea is the ²²²Rn activity (Bq m^-3) of seawater end-member, F_sea is the ²²²Rn flux via sediment diffusion (Bq m^-2 d^-1), ²²⁶Ra_sw is the ²²⁶Ra concentration in surface water, and A is the inundated area (m²).

Similar to the ²²²Rn calculation, carbon outwelling (F_outwelling, mmol m^-2 d^-1) from intertidal creeks was estimated as follows:

where C_sw is the concentration of carbon species in surface water (mmol L^-1) and C_sea is the corresponding seawater endmember of the carbon species (mmol L^-1).

Greenhouse gas emissions at the water-air interface were calculated from a bulk flux equation (Wanninkhof, 2014); therefore, greenhouse gas emissions (F_emissions, mmol m^-2 d^-1), including CO₂ and CH₄, from creek water were estimated as follows:

where C_sw is the greenhouse gas concentration in surface water (mmol L^-1), C_air is the greenhouse gas concentration in air (mmol L^-1), and k is the gas transfer velocity (m d^-1), which was the mean value derived from three gas transfer models (Borges et al., 2004; Ho et al., 2016; Rosentreter et al., 2017), α is the solubility coefficient of greenhouse gas. Uncertainties regarding the ²²²Rn mass balance model and carbon fluxes are estimated based on the basic rules of error propagation.

3 Results and Discussion

3.1 Surface Water and Porewater Observations

During the surface water observation, temperature and salinity were found with spatial gradients, whereas DO and pH were relatively stable (Figure 2 and Table 1). The surface water temperature increased from downstream (20.4°C) to upstream (28.7°C) while the salinity showed a contrasting trend decreasing from 13.7 to 0.5. Surface water DO and pH were irregularly distributed in ranges of 54–107% (4.7–8.6 mg L^-1) (mean: 94 ± 10%, 7.6 ± 0.7 mg L^-1) and 7.1–8.2 (mean: 7.9 ± 0.3), respectively, and the lowest pH were measured at upstream of creeks. ²²²Rn, carbon, and greenhouse gases showed large spatial heterogeneity, indicating the necessity for spatial investigation (Figure 3). Surface water parameters varied over a range of 10–521 (mean: 81 ± 103) Bq m^-3 for ²²²Rn, 1.54–7.90 (mean: 2.31 ± 1.36) mmol L^-1 for DIC, 0.23–0.79 (mean: 0.45 ± 0.14) mmol L^-1 for DOC, 29–179 (mean: 51 ± 32) μmol L^-1 for CO₂ and 94–939 (mean: 235 ± 140) nmol L^-1 for CH₄. Carbon species in surface water were dominated by DIC with various DOC proportions (12%–26%) and negligible greenhouse gases (Figure 4).

Figure 2 Spatial distributions of (A) temperature, (B) salinity, (C) DO and (D) pH in surface water and porewater.

Table 1 Summary of surface water observations.

Figure 3 Spatial distributions of (A) ²²²Rn, (B) DIC, (C) DOC, (D) CO2 and (E) CH₄ in surface water and porewater.

Figure 4 Ternary diagram illustrating the percentage of different carbon species [DIC, DOC and greenhouse gases (GHGs)] in surface water and porewater.

All hydrological parameters in porewater samples showed spatial heterogeneity (Figures 2, 3 and Table 2). Temperature, salinity, DO and pH changed from 22.6 to 26.3°C, 4.7 to 11.7, 0.5 to 58.6% (0.03 to 4.73 mg L^-1) and 7.04 to 7.54, with mean values of 24.6 ± 1.2°C, 8.71 ± 2.46, 13.8 ± 19.3% (1.2 ± 1.5 mg L^-1) and 7.32 ± 0.16, respectively. Porewater ²²²Rn activities varied from 1.01×10³ Bq m^-3 to 4.91×10³ Bq m^-3 with the mean value of (1.95 ± 2.02)×10³ Bq m^-3, which was approximately 24-fold higher than that in surface water. Carbon and greenhouse gases displayed considerable variability in porewater. As expected, DIC (range: 5.6–15.4 mmol L^-1, mean: 10.1 ± 3.0 mmol L^-1), DOC (range: 0.28–1.78 mmol L^-1, mean: 0.85 ± 0.41 mmol L^-1), CO₂ (range: 325–1280 μmol L^-1, mean: 709 ± 277 μmol L^-1) and CH₄ (range: 551–138400 nmol L^-1, mean: 6580 ± 4510 nmol L^-1) were highly enriched in porewater, which were approximately 4.5, 1.9, 14.2 and 28.1 times their respective concentrations in surface water. Similarly, in porewater, the major carbon species was also DIC, while DOC and greenhouse gases were minor components (Figure 4). This is because sulfate reduction coupled to pyrite formation effectively convert sediment organic carbon into bicarbonate (the main component of DIC) (Reithmaier et al., 2021).

Table 2 Summary of porewater observations.

3.2 Source Identification of Organic Carbon in Sediments and Porewater

According to different photosynthetic processes, plants can be divided into C3 and C4 plants, with distinct differences in the proportion of ¹³C isotopes. Generally, the δ¹³C values of C3 plants (range from -34‰ to -23‰) were more negative than those of C4 plants (range from -17‰ to -9‰) (Chmura and Aharon, 1995). In the Andong Shoal, local saltmarsh species, Scirpus mariqueter, Suaeda glauca, and Phragmites australis, were typical C3 plants with δ¹³C in range from -29‰ to -27‰, but the C4 plant Spartina alterniflora had a much higher δ¹³C of approximately -14‰ (Table 3 and Figure 5). For each plant species, δ¹³C values were relatively constant for various C/N ratios in the different organs (Figure 5).

Table 3 C/N molar ratio and δ¹³C value of vegetations in Andong Shoal.

Figure 5 Stable carbon isotope of organic carbon in surface water, porewater, sediment and vegetations (including Scirpus mariqueter, Spartina alterniflora, Suaeda glauca and Phragmites australis), and corresponding C/N molar ratio.

Combining organic δ¹³C values with C/N ratios in sediments and porewater can trace the source of organic carbon (Meyers, 1994). In sediment samples, results of δ¹³C (range from -25.0‰ to -23.8‰) and C/N ratio (range from 9.79 to 11.42) implied that the C3 plant Scirpus mariqueter was the major source of sediment organic carbon (Figure 5 and Tables 3, 4). A low C/N ratio (<10) may indicate that organic carbon was provided by lake or marine algae (Meyers, 1994). While lake algae would not be the source of organic carbon as no direct connection with lake ecosystems, marine algae can be a potential source because of frequent algal blooms around Hangzhou Bay (Liu et al., 2013). Sediment organic carbon was not influenced by the invasion of Spartina alterniflora, because of the low density in our study region. Furthermore, in the porewater samples, δ¹³C values of DOC were relatively constant at -26‰, but C/N ratios varied from 22.28 to 79.48 (Table 4). Here, we suggest that porewater-derived DOC flux was mainly provided by the biomass of Scirpus mariqueter due to approximate δ¹³C value (Figure 5).

Table 4 C/N molar ratio and δ¹³C value in sediment, surface water and porewater samples.

3.3 ²²²Rn-Based Porewater Exchange Rate and Associated Carbon and Greenhouse Gas Fluxes

To access the ²²²Rn fluxes via porewater exchange in the saltmarsh, all ²²²Rn sources and sinks were quantified (Figure 6). According to the ²²²Rn mass balance model (Equation 1), the ²²²Rn flux via porewater exchange was 196 ± 87 (Bq m^-2 d^-1), which accounted for 64% of the total ²²²Rn sources. In contrast, ²²²Rn fluxes (Bq m^-2 d^-1) via influx during flood tide, sediment diffusion, and ²²⁶Ra decay accounted for 22%, 13%, and 0.1% of ²²²Rn sources, respectively. Similar results of sediment diffusion and ²²⁶Ra decay were found in other coastal wetlands (Santos et al., 2019; Chen et al., 2021a; Chen et al., 2021b; Wu et al., 2021). In terms of the ²²²Rn sinks, outflux during the ebb tide, atmospheric evasion, and ²²²Rn decay accounted for 55%, 41%, and 4%, respectively. ²²⁶Ra decay and ²²²Rn decay were minor components in the ²²²Rn mass balance model and were negligible because of the relatively low percentage of ²²²Rn sources or sinks.

Figure 6 The ²²²Rn sources and sinks (Bq m^-2 d^-1) in Andong Shoal.

Determining the porewater endmember is the key step in estimating the porewater exchange rate, which has been considered a major source of uncertainty (Moore and Arnold, 1996). As the large spatial variation of natural tracer concentrations in aquifers (Peterson et al., 2009), collecting numbers of representative sample can help deal with uncertainty (Correa et al., 2021). In this study, to reduce the uncertainty caused by porewater endmember, we conducted a spatial investigation of porewater samples (n=9, Figure 1). Here, the porewater endmember was defined as the difference between the median porewater concentration and the median concentration of surface water at the creek mouth (Taillardat et al., 2018). Hence, the radon-derived porewater exchange rate was estimated to be 5.60 ± 2.78 cm d^-1 using ²²²Rn flux via porewater exchange divided by the porewater ²²²Rn endmember. This porewater exchange rate is in the range (3.4–12 cm d^-1) of other saltmarsh studies, as summarized by Liu et al. (2021).

Porewater exchange drives the transport of carbon species from the sediment to surface water. This can be proven by the significant positive correlations (Figure 7) between ²²²Rn and DIC (R^{2 =}0.49, p<0.001), DOC (R^{2 =}0.27, p<0.001), CO₂ (R^{2 =}0.60, p<0.001), and CH₄ (R^{2 =}0.62, p<0.001) in surface water and higher concentrations of ²²²Rn and carbon species in porewater than those in surface water (Figure 7). Therefore, we used the difference in median carbon or greenhouse gas values between porewater and surface water as the porewater endmember. By multiplying the porewater exchange rate with the corresponding carbon and greenhouse gas concentrations of porewater endmembers, the porewater-derived carbon and greenhouse gas fluxes (mmol m^-2 d^-1) were estimated to be 447 ± 227 (DIC), 26 ± 20 (DOC), 40 ± 21 (CO₂), and 0.25 ± 0.13 (CH₄) (Table 5). Most of the porewater-derived carbon flux was contributed by DIC (~90%) rather than DOC or greenhouse gases. Similar results for DIC, DOC, and CO₂ were obtained from a saltmarsh in the USA (Correa et al., 2021). However, porewater-derived carbon flux is mainly sourced from DOC in some other saltmarshes (Santos et al., 2019; Chen et al., 2022). This may be due to their dominant species having higher net primary productivity, leading to the rapid accumulation of organic carbon that can be enriched in porewater (Chen et al., 2022).

Figure 7 Correlations of DIC, DOC, CO₂ and CH₄ with ²²²Rn for surface water samples. Porewater samples are included for comparison.

Table 5 Carbon outwelling and greenhouse gas emissions (mmol m^-2 d^-1) in Andong Shoal.

3.4 Implications of Porewater–Derived Carbon Outwelling and Greenhouse Gas Emissions on Saltmarsh Blue Carbon Budget

3.4.1 Carbon Outwelling and Greenhouse Gas Emissions

The outwelling fluxes of DIC, DOC, CO₂ and CH₄ were estimated to be 1200 ± 61, 115 ± 70, 36.5 ± 0.5, and 0.13 ± 0.01 (mmol m^-2 d^-1) (Table 5), indicating that tidal creeks were net exporters of DIC, DOC, and greenhouse gases. Carbon outwelling was dominated by DIC (~90%) with minor contributions from DOC and greenhouse gases, providing further evidence that carbon outwelling flux is generally dominated by DIC in saltmarshes (Santos et al., 2021). The DIC outwelling flux (1200 mmol m^-2 d^-1) was very close to that of the Chongming Dongtan saltmarsh (Yangtze River Estuary, China) (1050 mmol m^-2 d^-1) in the nearby study area investigated by Liu et al. (2021). However, this exceeded the outwelling flux range (9–680 mmol m^-2 d^-1) in other study areas (Neubauer and Anderson, 2003; Wang and Cai, 2004; Wang et al., 2016; Chu et al., 2018; Czapla et al., 2020; Chen et al., 2022), which may be due to the macrotidal environment at our study site.

CO₂ and CH₄ emission fluxes through the water-air interface were estimated to be 54.63 ± 0.45 and 0.19 ± 0.01 (mmol m^-2 d^-1) (Table 5), implying that tidal creeks of saltmarsh are greenhouse gas sources for atmosphere. The CO₂ emission flux (54 mmol m^-2 d^-1) was within the emission flux range (2–288 mmol m^-2 d^-1) reported in previous studies (Neubauer and Anderson, 2003; Wang and Cai, 2004; Chmura et al., 2016; Chen et al., 2022). Meanwhile, the CH₄ emission rate (0.19 mmol m^-2 d^-1) in our study area (multi-species saltmarsh) was lower than the emission rate range (0.23–1.29 mmol m^-2 d^-1) of other saltmarshes covered by Spartina patens (Chmura et al., 2016; Chen et al., 2022). Methylamines released by decaying Spartina alterniflora (Wang and Lee, 1994) can be converted to CH₄ via microorganisms (Yuan et al., 2019; Seyfferth et al., 2020) and stored in the sediment.

3.4.2 Role of Porewater-Derived Carbon Fluxes

Organic carbon from in situ primary production can be buried in sediments because of the accumulation of detritus and roots (Alongi, 2020; Correa et al., 2021). As carbon burial is a function of mitigating climate change (Duarte et al., 2013; Wang et al., 2021), many previous studies relating to saltmarshes have focused on carbon burial rates (Herrmann et al., 2015; Najjar et al., 2018). The carbon burial rate in Andong Shoal was 140 g m^-2 yr^-1 (Xia et al., 2019). However, we found that part of the sediment carbon could be flushed out via porewater exchange, which may lead to an important revision of the saltmarsh blue carbon budget.

To approach the contribution of porewater exchange to the saltmarsh blue carbon budget, we constructed a conceptual model of major carbon flows (Figure 8). Some of the buried organic carbon can be converted to DIC by sulfate/Fe-oxide reduction (Santos et al., 2019; Santos et al., 2021; Zhu et al., 2021), whereas DOC species are released from biomass. While porewater exchange contributed to 60% of DIC and 36% of DOC outwelling, the DIC outwelling flux was 10-fold that of DOC. Our estimated DIC flux via porewater exchange and DIC outwelling were 1.2-fold and 3.2-fold of carbon burial, respectively. These results were similar to those of a recent investigation of Chongming Dongtan saltmarsh (Liu et al., 2021), where DIC export was 3-fold greater than local carbon burial. Overall, the carbon burial rate (9.42×10⁵ mol d^-1) accounted for 74% of the porewater-related carbon fluxes (1.27×10⁶ mol d^-1) and 28% of the carbon outwelling (3.34×10⁶ mol d^-1). Hence, porewater-derived carbon outwelling can be considered a mechanism for long-term carbon sink because bicarbonate (the dominant species in DIC) can remain in the ocean for 100,000 yr under a relatively stable pH circumstance (Santos et al., 2019; Middelburg et al., 2020; Xin et al., 2022; Yau et al., 2022).

Figure 8 Conceptual model of major carbon flows (including carbon burial, porewater exchange, carbon outwelling and GHG emissions, mol d^-1) in Andong Shoal.

Greenhouse gases were minor components of porewater-derived carbon fluxes compared with DIC fluxes (Figure 8). The CO₂ (9.92×10⁴ mol d^-1) and CH₄ (6.06×10² mol d^-1) fluxes via porewater exchange contributed 75% and 100% of those fluxes in atmospheric evasion, respectively. Although the CO₂ and CH₄ fluxes were at least one order of magnitude lower than the carbon burial rate, their greenhouse effects cannot be ignored. Converting CH₄ fluxes into CO₂ equivalents by global warming potential values of 96 for emission time frames of 20 yr (Alvarez et al., 2018), and converting molar units to mass units. Here, the CO₂-equivalent greenhouse gas emissions would be 6.7 t CO₂-C d^-1, while total sediment carbon burial would be 41.4 t CO₂-C d^-1 in Andong Shoal. Therefore, porewater-derived greenhouse gas emissions may offset 16% of sediment carbon burial.

4 Conclusions

In this study, based on a spatial survey of porewater, surface water, sediment, and saltmarsh plants in a subtropical multi-species saltmarsh, we draw the following conclusions:

(1) The stable carbon isotope (δ¹³C) and C/N ratio suggest that the dominant C3 species Scirpus mariqueter, is the main organic carbon source for the sediment and water column when study area is invaded by C4 species Spartina alterniflora.

(2) There was 5.60 ± 2.78 cm d^-1 of ²²²Rn-based porewater exchange rate, which implicated porewater-derived DIC, DOC CO₂ and CH₄ fluxes (mmol m^-2 d^-1) at 447 ± 227, 26 ± 20, 40 ± 21 and 0.25 ± 0.13, respectively. Porewater-derived DIC and DOC fluxes supported 60% and 36% of the corresponding species in carbon outwelling.

(3) Combining our results (porewater exchange, carbon outwelling, and greenhouse gas emissions) with literature data (i.e., carbon burial), porewater-derived DIC flux and DIC outwelling flux were 1.2-fold and 3.2-fold that of carbon burial, respectively. In addition to saltmarsh carbon burial, the DIC input to the ocean can be an important carbon sink because DIC can remain for a long duration.

(4) Although CO₂ and CH₄ were minor components in carbon pathways compared with DIC, their water-air emissions contributed by porewater carbon can offset 16% of the saltmarsh carbon sequester.

Overall, we highlight the importance of porewater exchange-related carbon outwelling as a long-term carbon sink in multi-species saltmarshes and the potential fate of atmospheric carbon fixed by saltmarsh vegetation. These provide a scientific basis for the protection and restoration of saltmarshes in the context of global climate change. The seasonal change and the organic carbon lability in saltmarshes deserve further studies because of their influence on quantification of blue carbon flux and evaluation of potential carbon sink.

Data Availability Statement

The original contributions presented in the study are included in the article/supplementary material. Further inquiries can be directed to the corresponding authors.

Author Contributions

PZ, XC, and LL designed the study; XC, YZ, QZ, XW, HZ, and LQ conducted the field work; PZ and XC performed the experiments and analyzed the data. PZ wrote the manuscript with contributions from all authors. All authors read and approved the final manuscript.

Funding

This research was supported by the Zhejiang Provincial Natural Science Foundation of China (LQ21D060005), Natural Science Foundation of China (42006152) and China Postdoctoral Science Foundation (2020M681931).

Conflict of Interest

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Publisher’s Note

All claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. Any product that may be evaluated in this article, or claim that may be made by its manufacturer, is not guaranteed or endorsed by the publisher.

Acknowledgments

We would like to thank Danping Huang for her kind assistance in the laboratory.

References